Phenols contaminated soils

Fig. 20. A typical GC-MS trace of a phenol contaminated soil sample, Bitterfeld, Germany (after [254] with permission). Chlorophenols were extracted using ASE-SPME upper chromatogram, procedure B lower chromatogram, ASE conditions of water, 150°C, 15 min. Peak identifications (1) 2-chlorophenol, (2) 2,4-dichlorophenol, (3) 4-chlorophenol, (4) 4-chloro-3-methylphenol, (5) 2,3,5-trichlorophenol, (6) 2,4,6-trichlorophenol, (7) 2,3,4-trichlo-rophenol, (8) 2,3,4,6-tetrachlorophenol, (9) pentachlorophenol... 

Luo QS, Wang H, Zhang XH, Fan XY, Qian Y. (2006). In situ bioelectrokinetic remediation of phenol-contaminated soil by use of an electrode matrix and a rotational operation... 

Luo Q, Zhang X, Wang H, Qian Y. (2005). The use of non-uniform electrokinetics to enhance in situ bioremediation of phenol-contaminated soil. Journal of Hazardous Materials B121 187-194. 

Figure 213. The distribution of electric potential difference across the soil matrix in a sandbox scale remediation of phenol-contaminated soil by the EK-Fenton process after 20 days of reaction.

Chen YS. (2002). Treatment of Phenol-Contaminated Soils by Combined Electrokinetic-Fenton Process. MS Thesis, National Sun Yat-Sen University, Kaohsiung, Taiwan (in Chinese). 

Yang GCC, Lai WH. (1997). Chemical oxidation treatment of phenol-contaminated soil by Fenton process. 1997 Extended Abstracts for the ACS Special Symposium on Emerging Technologies in Hazardous Waste Management IX, September 15-17, 1997, Pittsburgh, PA, p. 107. 

Yang GCC, Long YW. (1998). Treatment of phenol-contaminated soil by electrokinetics-Fenton process. ACS Special Symposium on Emerging Technologies in Hazardous Waste Management X, Book of Abstracts, 21 ACS National Meeting, August 23-27, 1998, Boston, MA. 

Yang GCC, Long YW. (1999a). Treatment of phenol contaminated soil by in-situ electrokinetic remediation and Fenton-like process. Proceedings of the Second Symposium on Heavy Metals in the Environment and Electromigration Applied to Soil Remediation, July 7-9,1999, Lyngby, Denmark, pp. 65-70. 

Hilarides and others (1994) investigated the destruction of TCDD on artificially contaminated soils using °Co y radiation. It appeared that TCDD underwent stepwise reduction dechlorination from tetra- to tri-, then di- to chlorodioxin, and then to presumably nonchlorinated dioxins and phenols. The investigators discovered that the greatest amount of TCDD destruction (92%) occurred when soils were amended with 25% water and 2% nonionic surfactant [alkoxylated fatty alcohol (Plurafac RA-40)]. Replicate experiments conducted without the surfactant lowered the rate of TCDD destruction. 

Kahru, A., Maloverjan, A., Sillak, H. Pollumaa, L. 2002. The toxicity and fate of phenolic pollutants in the contaminated soils associated with the oil-shale industry. Environmental Science and Pollution Research International (Special Issue), 1, 27-33. 

Up to 47 mg/kg of CP-transformation products such as o- and />-hydroxylated phenols (Knuutinen et al., 1990), as well as chloroanisoles such as 2,3,4,6-TeCA and PCA (Palm et al., 1991), have often been found in CP-contaminated soils. An additional route for contamination is the CP-treated utility poles and railway ties that contaminate nearby environments via runoff and leaching (Wan, 1992). 

If the skin or the clothes are contaminated with phenols, the soiled clothes should be removed at once, and the skin flushed with warm water and washed with dilute alcohol. When working with phenols, goggles should always be worn. Cresols are similarly poisonous, but are less-toxic than phenol. Napthols are much less irritant and toxic... 

Figure 4 shows the results of the extraction of water (figure 4a) and dry and wetted soil (figure 4b and 4c, respectively) using pure carbon dioxide, carbon dioxide with 2 mol % benzene, and carbon dioxide with 2 mol % methanol at 15 MPa and 298 K. For the extraction of dry contaminated soil, the distribution coefficient of phenol between the soil and pure carbon dioxide was 0.35, as shown in Figure 4b. The presence of benzene increased the distribution coefficient almost 100 %, while the presence of methanol resulted in the removal of essentially all of the phenol from the soil (within experimental accuracy, K-values > 7 correspond to almost complete removal). For the extraction of wetted soil (10 wt.% water )with pure carbon dioxide the distribution coefficient of phenol was again 0.35. The effect of the entrainers on this system, however.

Example 7.2 Shake-Flask Extraction of Phenols from Contaminated Soil... 

Figure 7.6 Results obtained for the shake-flask extraction of various phenols from contaminated soil and Celite A, phenol B, 3-cresol C, 4-ethylphenol D, 1-naphthol , Celite . soil [2] (cf. DQ 7.4).

UV spectra of soil B present a marked shoulder at 225 nm and a significant absorbance up to 350 nm. Small shoulders are observed around 250 nm and 270-280 nm. These particularities are characteristic of industrial pollutants such as phenols, which can be found in PAH-contaminated soils and compounds belonging to the PAH family. Moreover, the residual pollution is more important in soil B. 

DEFRA and Environment Agency (In prep) CLR 10 GV8 Guideline values for phenol contamination in soils. 

It is now obvious that atmospheric transport of persistent toxic organic substances is the major pathway between ecosystems. For dioxin, volatilization of residues from contaminated soils was first noted as a concern at Seveso, Italy (4). The National Research Council of Canada reported that atmospheric emissions were the major source of chlorinated dioxins in the Canadian environment (5). A recent Ontario report estimates that from 8 10 kg of 2,3,7,8 -TCDD equivalents enter the Ontario environment annually from combustion of municipal refuse and sewage sludge and that all other combustion sources contribute from 20 -50 kg annually (6). The only other major source considered was from the use and disposal of chlorinated phenols. 

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